Steal the rain: Interception loses and rainfall partitioning by a broad‐leaf and a fine‐leaf woody encroaching species in a southern African semi‐arid savanna

Abstract Woody plant encroachment (WPE) has been found to alter ecosystem functioning and services in savannas. In rain‐limited savannas, increasing woody cover can reduce streamflow and groundwater by altering evapotranspiration rates and rainfall partitioning, but the ecological relevance of this impact is not well known. This study quantified the altered partitioning of rainfall by two woody plant structural types (fine‐ and broad‐leaved trees) across a gradient of encroachment in a semi‐arid savanna in South Africa. Averaged across both plant functional types, loss of rainfall through canopy interception and subsequent evaporation roughly doubled (from 20.5% to 43.6% of total rainfall) with a roughly 13‐fold increase in woody cover (from 2.4 to 31.4 m2/ha tree basal cover). Spatial partitioning changes comprised fourfold increases in stemflow (from 0.8% to 3.9% of total rainfall) and a decline in throughfall proportion of about two‐fifths (from 80.2% to 47.3% of total rainfall). Changes in partitioning were dependent on plant functional type; rainfall interception by the fine‐leaved multi‐stemmed shrub Dichrostachys cinerea was almost double that of the broad‐leaved tree Terminalia sericea at the highest levels of woody encroachment (i.e., 49.7% vs. 29.1% of total rainfall intercepted at tree basal area of 31.4 m2/ha). Partitioning was also dependent on rainfall characteristics, with the proportion of rainfall intercepted inversely related to rainfall event size and intensity. Therefore, increasing tree cover in African grassy ecosystems reduces the amount of canopy throughfall, especially beneath canopies of fine‐leaved species in smaller rainfall events. Rainfall interception traits may thus confer a selective advantage, especially for fine‐leaved woody plant species in semi‐arid savannas.


| INTRODUC TI ON
Savannas are characterized by discontinuous tree canopy in a continuous grass layer and cover about 20% of the Earth's and over 50% of Africa's land surface area (Scholes & Archer, 1997;Wang et al., 2009). Savannas are experiencing significant increases in woody plant encroachment-where indigenous woody cover is increasing (Stevens et al., 2017;Venter et al., 2018). The continued increase in woody cover within non-forested systems threatens biodiversity and alters the structure and function of savannas and the ecosystem services they provide (de Klerk, 2004;Eldridge et al., 2011;Meik et al., 2002). The increased woody cover shades out the grassy layer, reducing grass biomass and hence forage availability (Belay & Moe, 2015;Charles-Dominique et al., 2018;Randle et al., 2018).
In water-limited systems, woody encroachment impacts the ecosystem hydrology by reducing above-and below-ground water availability through increasing evapotranspiration (Archer, 2010;Grygoruk et al., 2014;Scott et al., 2006;Wang et al., 2018) when deeper-rooted trees access deeper soil layers resulting in drying the soil during transpiration (Scott et al., 2006). High levels of encroachment also cause water loss via evaporation through canopy interception, where rainfall landing on the leaves of a tree canopy remains on the leaves and gets evaporated (Dohnal et al., 2014;Honda & Durigan, 2016). The partition of rainfall into interception, throughfall, and stemflow has been extensively quantified and documented in forest systems, however, similar studies are still lacking in savanna systems, especially in Africa (Magliano et al., 2019). In forests, canopy interception losses have been shown to reduce as much as 10%-50% of rainfall reaching the ground, with this amount varying with forest characteristics and climate (Carlyle-Moses & Gash, 2011;Roth et al., 2007). Similarly, in arid shrublands, as much as 9%-25% of rainfall can be lost to interception by vegetation canopies (Magliano et al., 2019;Návar et al., 1999;Zhang et al., 2015Zhang et al., , 2017). Yet, we cannot generalize findings from other biomes to savanna ecosystems due to differences in dominant plant functional types and the differences in the stem and canopy architectures of the trees. Forest trees, for example, are taller with wider canopy diameter for a given basal area and have higher specific leaf area (Archibald & Bond, 2003;Ratnam et al., 2011). This, therefore, remains a significant gap in savannas, especially African savannas, as it is not well documented how much canopy interception occurs generally and or how this component of the water cycle shifts with woody encroachment (Honda & Durigan, 2016;Savenije, 2004).
The relationship between canopy interception and encroachment might also be altered by the type of rainfall. A small and less intense rainfall event is more likely to have more rain intercepted by the canopy and evaporated back into the atmosphere.
Rainfall in semi-arid savannas is characterized by a few large rainfall events and several small rainfall events while mesic savannas are characterized by a few small rainfall events but many large rainfall events (Pilgrim et al., 1988). If this holds true, encroached arid and semi-arid savannas that receive relatively small rainfall events will experience more significant losses of rainfall through interception.
The architecture of trees is also likely to be a crucial factor that shapes how much rainfall is lost to interception. In Southern African semi-arid savanna systems, where woody encroachment is prevalent (Stevens et al., 2017), encroachment is dominated by two plant functional types; thorny fine-leaved leguminous shrubs such as Dichrostachys cinerea, Vachellia, and Senegalia species, and by broad-leaved trees such as Terminalia sericea and Combretum species (Ben-Shahar, 1992;Roques et al., 2001). Savanna broad-leaf trees are shorter than forest trees but are taller and have wider canopies than fine-leaved species (Moncrieff et al., 2014). Fine-leaved species on the other hand are relatively shorter and shrubby with wide and round canopies that are much closer to the ground (Moncrieff et al., 2014). Therefore, the architectural differences between these functional types (Randle et al., 2018) may result in differences in rainfall partitioning, as previous studies show architectural differences lead to distinct ecosystem impacts when their cover increases (Belay & Moe, 2015;Moncrieff et al., 2014;Osborne et al., 2018;Randle et al., 2018;Zizka et al., 2014).
To address this gap, we examined how the partitioning of rainfall changed across the gradient of woody plant encroachment in a semiarid African savanna. We investigated how this relationship was modified by (i) plant functional types (fine-leaf D. cinerea vs. broadleaf T. sericea) and (ii) rainfall characteristics (size and intensity).

| Study area
This study was located at Wits Rural Facility (WRF; 24°31′S; 31°06′ E), a 350-ha research station of the University of the Witwatersrand, in the Lowveld savanna within the Limpopo Province of South Africa.

| Sampling procedure
To investigate the influence of woody plant encroachment on rainfall partitioning, we established three 5 × 5 m plots per species across a gradient of woody encroachment with each plot replicated three times. This was repeated for two species (Dichrostachys cinerea and Terminalia sericea) ( Figure 1, and see Randle et al., 2018, for a detailed description of these two species). Three levels of encroachment were selected: low, medium, and high. The levels of encroachment were initially characterized by stem counts in the 5 × 5 m plots. Low encroachment plots were represented by 1-2 individual trees, medium by 5-6 individual trees, and high by more than 10 individual trees (Figure 1). Between the two species, D. cinerea has lots of stems and T. sericea does not, therefore, to standardize, stems further than 30 cm apart were counted as separate trees. To avoid influence by other tree species, we only selected plots that exclusively contained the study species of interest (D. cinerea and T. sericea). Every treatment (species × encroachment level) was replicated three times with three 25 m 2 plots located between 0.5 and 2 km from each other. No plot was located more than 2 km apart to ensure similar rainfall events and soil conditions. For multi-stemmed trees, we defined individual trees as single stems coming from the ground more than 30 cm apart.

| Measurements of vegetation characteristics
At the beginning of the study, each 25 m 2 plot was surveyed to characterize vegetation. For each tree, we measured height, stem diameter (at 0.5 m height), stem density (number of stems per plot), and canopy cover (the percentage of ground area shaded by overhead foliage). The canopy cover was quantified using a Cl 110 Plant F I G U R E 1 The experimental design to measure gross precipitation (2 × rain gauges in the open spaces outside each plot), throughfall (4 × rain gauges inside each plot), and stemflow (collected using buckets attached to stems) across a gradient of woody encroachment (low, medium, and high) for Dichrostachys cinerea and Terminalia sericea. The two pictures represent a highly encroached plot for each of the two species.
Canopy Imager (https://cid-inc.com/) in the form of leaf area index (LAI). Measurements were taken by extending the arm inside the plot every 2.5 m along the perimeter of the plot, adding to a total of 8 points measured inside a 5 m × 5 m plot. Due to the wide field of view of the fish-eye lens, eight measurements covered the entire area of the plot. Canopy cover was done during summer for all plots to reduce seasonal bias. Dense stands (highly encroached) of D. cinerea had multiple thin stems with a high canopy cover (Table S1; Figure S1), and dense stands (highly encroached) of T. sericea on the other hand were characterized by few, thick stems with a lower LAI than D. cinerea (Table S1; Figure S1). Tree basal area (TBA) was calculated for each plot using the formula: where DBH is the diameter (m 2 ) of each stem within the plot at breast height and ha is the area of the plot.

| Measurements of rainfall partitioning and rainfall characteristics
The quantification of gross precipitation and rainfall partitioning into stemflow, throughfall, and interception was done for each plot (9 plots per species) during the rainy season between November and March of the years 2019-2020 and 2020-2021 when the trees were in full canopy. A rainfall event was defined as a measurable amount of rainfall separated from the previous or the next rainfall input by the time required for the foliage and trunks to dry (Krämer & Hölscher, 2009). In our study site, the foliage and trunk dried between 3 and 5 h, so each rainfall event was considered a separate event after 5 h had passed. In each plot, gross precipitation (the total amount of rain that falls on the ground in the open) was quantified using two rain gauges installed in open spaces ( Figure 1). Each rain gauge had a catchment area of 133 cm 2 and was installed at a height of 0.5 m aboveground. The amount of water collected in the rain gauge was measured using a measuring cylinder and then emptied after each rainfall event. The rain gauges for measuring throughfall and the buckets for measuring stemflow were coated with oil to avoid evaporation of the collected water. The duration of each rainfall event was obtained from a tipping bucket rain gauge installed in between the plots to be able to calculate rainfall intensity later.
Regular inspections and maintenance work was done between rainfall events to ensure that all rain gauges were in place and that no collars were broken.
Rainfall data were partitioned into throughfall, stemflow, and interception. To get a value equivalent to the standard mm of rainfall, each rainfall partition was calculated as per unit area (Lm − 2 ). The average gross precipitation from the two rain gauges installed around each plot (Figure 1) was calculated as: To measure throughfall in each plot, four rain gauges were installed beneath tree canopies ( Figure 1). Throughfall rain gauges were placed at a 2 m distance from the nearest plot corner (Figure 1), and they were placed so they did not touch any stems or branches to avoid heavy run-off from the trunks (Rutter, 1963). The rain gauges' positions within the respective plots were kept fixed to capture the intensities of different rainfall events. Rainfall in each rain gauge was measured after each rainfall event using measuring cylinders. Plotlevel throughfall and throughfall proportion were calculated as: Stemflow was quantified using collars (made of polyurethane foam) with an internal diameter of approximately 5 cm which were attached around every stem within the plot at a height of ~0.5 m from the ground (Honda & Durigan, 2016;Krämer & Hölscher, 2009). The collars were sealed with silicone sealant ensuring that water leakages are avoided. Flexible tubes channeled the water into containers ( Figure 1). The total stemflow and proportion of stemflow measured per plot in each rainfall event were calculated as: The total amount of rainfall (net) and the proportion of rainfall reaching the ground in the plots were calculated as: Canopy interception and the proportion of interception for each rainfall event in each plot were calculated as:

| Characteristics of rainfall at the study site
A total of 45 rainfall events were recorded during the two growing seasons between 2019 and 2021. Mean annual rainfall was 389.8 mm and rain events ranged from 0.5 to 49.7 mm with an average of 8.4 mm across rainfall events ( Figure 2). Rainfall intensity (gross × duration) ranged from 0.1 to 8.2 mm/h with an (2) Gross rainfall Lm −2 = mean rainfall in the open catchment area of rain gauge (3) Throughfall Lm −2 = mean plot rainfall catchment area of rain gauge (4) Proportion throughfall P tf = Throughfall Gross rainfall total plot stemflow area of the plot (6) Proportion stemflow P sf = Stemflow Gross rainfall  (Barthiban et al., 2012). The 45 rainfall events were clustered into three rainfall classes: 31 (68.9%) fell into the 0-10 mm (low) rainfall class ( Table 1); 9 events (20.0%) and 5 events (11.1%) in the 10-20 mm (medium); and >20 mm (large) rainfall classes, respectively ( Table 1).
The large rainfall class contributed 169.3 mm which is 43.4% of the total rainfall recorded, followed by the medium class with 124.3 mm (31.9%), and lastly, the low class with 96.2 mm (24.7%) ( Table 1). The large class had the highest rainfall intensity (3.9 mm/h) ( Table 1). It was followed by the medium with 2.7 mm/h and the low rainfall class with 1.6 mm/h rainfall intensity ( Table 1). Even though all plots were located within a 2 km radius, a few rainfall events showed local spatial variation. Therefore, to reduce the effect of this on the analysis, we selected 40 of the 45 events with a coefficient of variation of less than 15%, as done by Honda and Durigan (2016). To determine the distributions of the three rainfall partitions (proportion throughfall, stemflow, and interception), we used the "gamlss.dist" R package which contains about 59 types of distributions grouped into four sets ("realAll," "realline," "realplus," and "real0to1"), which can be used for modeling a continuous response variable using generalized additive models for location scale and shape (GAMLSS) (Rigby & Stasinopoulos, 2005). The function "fitDist" was used to fit "realAll" (all the 51 gamlss.family continuous distributions defined on the real line (i.e., "realline" and the real positive line, i.e., "realplus")) and "real0to1" (all eight gamlss.

| Data analysis
family continuous distributions from 0 to 1) on each of the rainfall partitions. The final marginal distributions were ranked by their generalized Akaike information criterion (GAIC) (Rigby & Stasinopoulos, 2005). When comparing the fitted distributions, we found that a beta ("BE") distribution was consistently in the top 2 of the distributions that best represented the data (number 1 for Throughfall and number 2 for Stemflow and Interception) together with other distribution types such as the Skewed Normal type 2 ("SN2"), the Generalized Gamma ("GG"), and the Box-Cox Power Exponential "BCPEo" (See the Figure S2a for the BE fitting). We, therefore, ran Generalized mixed effects models using the "gamlss" R package with the top 3 distributions for each of the rainfall partitions, proportion throughfall (P tf ), stemflow (P sf ), and interception (P int ) in response to TBA, species, rainfall class, and rainfall intensity class. To account for variability across sites, we used "site" as a random effect. The general setup of the functions F I G U R E 2 Gross rainfall and rainfall intensity for 45 rainfall events in the study area during the growing seasons from 2019 to 2021.

TA B L E 1
Characteristics of rainfall within the study area during the sampling period. for P tf , P sf , and P int as response variables to treatments (TBA, species, rainfall class, and rainfall intensity) as fixed effects and site as a random effect was as follows:

Rain intensity range (mm/h)
To determine the best model that represented each of the rainfall partitions, we compared the models using their AIC scores and the distributions of the model residuals using Q-Q plots. The best-fitting model is represented by having the lowest AIC score (Wagenmakers et al., 2004). Again, we found that the beta (BE)-based models consistently fitted the data distribution in comparison with other models, being ranked first for P tf , second for P sf after the generalized beta type 1 (GB1), and second for P int after generalized gamma (GG). To maintain consistency and avoid bias, we, therefore, used the beta distribution throughout (see the Figure S2b for the fitting of the residuals for BE models). The significance level for all tests was assumed at p < .05. To predict the response variables from the model outputs, the "ggpredict" function within the "ggeffects" package was used. For simplicity, and for creating graphs, the predicted proportions (P tf , P sf , and P int ) were transformed into percentages (P tf %, P sf %, and P int %) of the gross by multiplying by 100.

| RE SULTS
Woody encroachment changes rainfall partitioning by increasing interception and stemflow. The amount of rainfall intercepted by the tree canopies increased across the gradient (TBA: 2.4-31.4m 2 /ha) of woody encroachment. At the lowest woody cover, 20.5% of the rainfall was intercepted while at the highest woody cover 43.6% of the rainfall was intercepted ( Figure 3). As tree basal area increased the amount of rainfall reaching the ground through stemflow increased from 0.8% at the lowest TBA to 3.9% at the highest TBA (Table S2; Figure 3). This, however, did not offset the increased losses from interception as throughfall declined from 80.2% at the lowest TBA to 47.3% at the highest TBA resulting in an overall 33.6% decrease in the amount of rainfall reaching the ground with woody encroachment (Table S2; Figure 3).
This interaction between woody encroachment and rainfall partitioning was further modified by plant functional types. Rainfall partitioning significantly differed between the two species (p < .05) (  (Figure 4).
The relationship between woody encroachment and rainfall partitioning was further influenced by rainfall size and intensity (Table S2). The amount of rainfall event had a negative effect on the proportion of rainfall lost through interception, where significantly less rainfall was lost to interception and more was gained from increased stemflow during large rainfall events (Figure 5). At the highest level of woody encroachment, interception loss decreased from 43.7% for D. cinerea and 24.4 for T. sericea when rainfall events were small (0-10 mm) to 23.4% and 11.3%, respectively, when the events were large (>20 mm) ( Figure 5). As a result, less rain, 51.2% for D. cinerea and 71.3% for T. sericea, reached the ground during low rainfall events (0-10 mm) compared to 68.1% for the former and 83% for the latter at high rainfall sizes (>20 mm) within the dense plots (31.4 m 2 / ha; Figure 5).
Similarly, rainfall intensity also significantly altered interception losses (p = .03; Table S2) where the percentage of rainfall reaching the ground increased as rainfall intensity increased due to a decline in rainfall interception (Table S2; Figures 5 and 6). At the highest woody cover, low rainfall intensities resulted in higher interception losses of 43.6 for D. cinerea and 27.2% for T. sericea, whereas high intensities resulted in lower (26.5% and 14.8%, respectively) interception losses ( Figure 6). Ultimately, less rainfall reached the ground (51.2% for D. cinerea and 71.3% for T. sericea) during less intense rainfall events (0-2.5 mm/h), in comparison to 64.3% and 81.3% for the respective species during more intense events (2.5-7.5 mm/h; Figure 6).

| D ISCUSS I ON AND CON CLUS I ON
Woody encroachment significantly changes rainfall partitioning by increasing interception loss and stemflow and reducing throughfall.
Based on this study, this results in approximately 44% of rainfall captured by woody canopies and evaporated back into the atmosphere at the highest levels of encroachment. This relationship is modified by the type of encroaching plants and the characteristics of the rainfall regime (size and intensity). About 9% less rain enters the soil when a system is encroached by a fine-leaved multi-stemmed shrub such as D. cinerea rather than a broad-leaved tree-like T. sericea.
Notably, this relationship is also impacted by rainfall characteristics and encroached areas where rainfall intensity and size are frequently large, experience less loss to interception than areas where the rainfall regime is characterized by frequent small rainfall events.
We showed that rainfall partitioning changed across a gradient of increasing tree basal area where the increased cover increased interception and stemflow and decreased throughfall. A study in a mesic savanna in Brazil also demonstrated that an increase in interception and stemflow and a decline in throughfall occurred as woody cover increased over an encroachment gradient (Honda (11) gamlss(y % mixed effects + random effects, data, family) & Durigan, 2016). The increase in canopy cover results in fewer gaps within and between tree canopies and increases the capacity for canopies to hold more water. The particular effectiveness of shrubs in channeling rainfall has also been shown where increases in stemflow occurred with an increase in the number of stems per unit area and a lower angle of stem insertion as seen in shrubs (Levia & Frost, 2003;Zhang et al., 2017). Moreover, the multistems of a shrub such as D. cinerea are vertically oriented, somewhat like an "inverted cone," and likely making them more efficient in funneling stemflow to the stem bases. This is in contrast to the single-stemmed morphology of taller trees, with branches ramifying in different directions from a certain height (Li et al., 2008;Martinez-Meza & Whitford, 1996;Zhang et al., 2015).
The sensitivity of rainfall partitioning to plant functional type is an essential element to understand when modeling the impacts of encroachment on rainfall. The difference in rainfall partitioning is likely driven by species-specific characteristics-from growth form, canopy architecture, stem orientation or angle, branching, and leaf traits such as shape, size, and angle (Crockford & Richardson, 2000;Levia & Frost, 2003;Pérez-Suárez et al., 2014). There is evidence that leaves that are held vertically allow greater light penetration (Falster & Westoby, 2003) and likewise more rain -but also that highly branched canopies result in higher interception (Li et al., 2016;Pflug et al., 2021). The position of leaves on the shoot -clustered at the tips or distributed along the stem -can also impact net throughfall. T. sericea is probably on the extreme end of the throughfall F I G U R E 3 The accumulation of rainfall partitioning into interception, throughfall, and stemflow in response to an increase in tree basal area (TBA) as per the predictions of the beta regression model.

F I G U R E 4
The accumulation of rainfall partitioning into interception, throughfall, and stemflow in response to an increase in tree basal area (TBA) for Dichrostachys cinerea and Terminalia sericea as per the predictions of the beta regression model. spectrum, having its broad leaves clustered in groups at the branch tips, which are also generally held more vertically, and with a fairly tall unbranched main stem which could tend to increase throughfall. By contrast, D. cinerea has a highly branched stem (multi-stem), with more lateral branches and leaves distributed throughout the branch length (Figure 1). The canopy is spheroid and deep with a relatively small crown-base height compared to T. sericea, therefore, adding more water-holding capacity (Belay & Moe, 2015;Martens et al., 2000;Randle et al., 2018). In addition, bipinnate leaves (fine leaves) have a high surface area-to-volume ratio allowing more surface area to retain water to evaporate back into the atmosphere (as shown in Figure 1). Consistent with this, Khan (1999) reported a F I G U R E 5 Rainfall partitioning into interception (a), stemflow (b), and throughfall (c) across a gradient of TBA by the two species and rainfall classes. The black curves represent the predicted values of each partition, and the upper and lower bands represent 95% confidence intervals (95% CI). These curves with 95% CI are fitted on the actual dataset (black dots on the scatter plots).
higher interception loss (21.77% vs. 12.72%) by a fine-leaf Vachellia tortilis when compared to a broad-leaf Colophospermum mopane in an arid zone in India.
The pattern of shifting rainfall partitioning across a woody gradient is not only altered by the dominant woody encroaching species but also depends on the characteristics of the rainfall regime where small and low-intensity rainfall events resulted in the highest rate of interception. With large rainfall size and intensity, tree canopies and stems quickly become saturated and the proportion of net rainfall increases (Carlyle-Moses, 2004;Pérez-Suárez et al., 2014;Zhang et al., 2015). Carlyle-Moses (2004) showed a similar pattern in a semi-arid system in northeast Mexico where there was an increase in F I G U R E 6 Rainfall partitioning into interception (a), throughfall (b), and stemflow (c) across a gradient of TBA by the two species and rainfall intensity. The black curves are the predicted values of each partition, and the upper and lower bands represent 95% confidence intervals (95% CI) from the beta regression model. These curves with 95% CI are fitted on the actual dataset (black dots on the scatter plots).
throughfall with an increase in rainfall size until the canopy reached saturation at 20 mm. A similar relationship with rainfall regime has been documented across regions and biomes where a decline in relative interception loss due to canopy saturation occurs across multiple species (Owens et al., 2006;Zhang et al., 2015). Another explanation that is beyond the scope of this study could be linked to an increase in wind speed during stormy high-intensity rainfall events where windy conditions reduce the size of water captured by tree canopies. This can also explain the observed high variability in the observed data, especially with D. cinerea, a shrub with relatively thinner stems that can be easily shaken by the wind.
In this study, we note that woody encroachment by D. cinerea and T. sericea results in less rainfall reaching the ground, especially at lower rainfall sizes and intensities. This is likely to be a generic result of encroaching species with comparable stem and leaf traits and canopy architecture. Differences emanating from tree branching ratios, length, branch angle, and leaf characteristics could lead to significant differences in the proportions of rainfall partitioning.
When comparing the two plant species, we conclude that the interception by fine-leaved D. cinerea is more pronounced than the broad-leaved T. sericea. Debushing programs that target the proliferation of encroaching species in arid regions should therefore prioritize controlling fine-leaved encroachers for optimum impact.
This has important implications for conservation and management not only in savanna systems but also in all open grasslands that are threatened by woody encroachment. A reduction of ~10% in water availability is significant, especially when viewed in light of future changes in rainfall (Al-Ansari et al., 2014;Milly et al., 2005). Reducing the size of water entering the ground will also have multiple interactive effects on other ecosystem services. For example, less water will result in less grass growth, which is already increasingly limited by increased shading driven by woody encroachment (Belay & Moe, 2015;Randle et al., 2018). Alternatively, the decrease in available water could make these encroaching trees more susceptible to drought and heat-related death (Case et al., 2019).
These results highlight an important consequence of increasing tree cover in grassy ecosystems and provide a valuable counter to the argument for increasing tree cover in grassy ecosystems as a tool to increase carbon sequestration (Bastin et al., 2019;Bond et al., 2019;Tear et al., 2021). We show that aside from reducing carbon grass biomass and biodiversity, high tree cover will also significantly reduce effective rainfall, especially in these semi-arid systems (Andersen & Steidl, 2019;Randle et al., 2018). In addition to the established differences in canopy interception with plant functional types, there is a need for exploring the role of individual tree characteristics such as canopy architecture and leaf traits in providing a selective advantage in arid and semi-arid savannas. This perspective could be a valuable line of inquiry in further studies on the drivers and consequences of woody plant encroachment.

ACK N OWLED G M ENTS
We extend our gratitude to Mr. Happy Mangena for assisting with data collection. We also thank Prof. Wayne Twine for his support during data collection at Wits Rural Facility.

FU N D I N G I N FO R M ATI O N
The study was funded by the SA-ICON Project (P1CGC00) under a PhD studentship and the Seamless Forecasting System Capability Development Project (P1DCM00) within the Council for Scientific and Industrial Research (CSIR). We also thank the University of Stellenbosch for supporting the study.

CO N FLI C T O F I NTER E S T S TATEM ENT
The authors declare no competing interests.

DATA AVA I L A B I L I T Y S TAT E M E N T
The rain partitioning experimental data can be found in the Dryad Digital Repository (DOI: https://doi.org/10.5061/dryad.mw6m9 061s).